Anthropogenic Contaminants - ACS Symposium Series (ACS

Chapter 6

Anthropogenic Contaminants Atmospheric Transport, Deposition, and Potential Effects on Terrestrial Ecosystems 1

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Downloaded by UNIV OF AUCKLAND on September 18, 2017 | http://pubs.acs.org Publication Date: February 4, 1992 | doi: 10.1021/bk-1992-0483.ch006

Thomas J. Moser , Jerry R. Barker , and David T. Tingey 1

ManTech Environmental Technology Inc., 200 SW 35th Street, Corvallis, OR 97333 Environmental Research Laboratory, U.S. Environmental Protection Agency, 200 SW 35th Street, Corvallis, OR 97333

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Through the processes of atmospheric transport and deposition, many anthropogenic contaminants such as industrial organics, pesticides, and trace metals have become widely distributed around the globe. Due to the phenomenon of long-range atmospheric transport, even the most remote areas of the planet are not out of range of contaminants emitted from distant anthropogenic sources. Many of these airborne contaminants are toxic and persistent, can bioaccumulate, and may remain biologically harmful for long periods of time. Although airborne contaminants are considered primarily a human health problem, there is increasing concern that they may have deleterious ecological consequences. When sensitive terrestrial plants and other biota experience chronic exposure to low concentrations of airborne toxic chemicals, sublethal effects may occur, with subsequent impacts on ecosystem structure and function. A large variety and quantity of contaminants are being released into the environment from point, area, and mobile anthropogenic sources. Once released, these contaminants may become widely dispersed via the fluid dynamics of surface waters and the atmosphere. The atmosphere is responsible for the long-range dissemination of contaminants over regional, hemispherical and global scales due to its dynamic nature and its ability to move contaminants rapidly. Through the processes of atmospheric transport and deposition, toxic chemicals have found their way to remote environments far from emission sources. Recent data strongly suggest that the enriched concentrations of several contaminants detected in the abiotic and biotic components of rural and remote environments are the result of long-range atmospheric transport from urban-industrial and agricultural sources (i-6). Many of these chemicals are toxic and persistent, can bioaccumulate, and may remain biologically active for long periods of time. 0097-6156/92/0483-0134$06.00/0 © 1992 American Chemical Society Dunnette and O'Brien; The Science of Global Change ACS Symposium Series; American Chemical Society: Washington, DC, 1992.


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An airborne pollutant can be broadly defined as any chemical occurring in the atmosphere in concentrations and exposure durations that may pose a threat to human health or the environment. This broad definition includes an array of chemicals ranging from the criteria pollutants (e.g., ozone, sulfur dioxide), which have resulted in well-documented biological effects at local and regional scales, to the greenhouse gases (e.g., methane, chlorofluorocarbons), with their implications for global warming and stratospheric ozone depletion. Another group of chemicals, often referred to as 'air toxics' or 'airborne contaminants', include a large number and variety of chemical species broadly categorized as industrial organics, agricultural pesticides, and trace metals and metalloids. These contaminants have strong anthropogenic emission sources and are known to be transported long distances (hundreds to thousands of kilometers) in the troposphere before being deposited into remote environments. The recent publication of the U.S. Environmental Protection Agency's Toxic Release Inventory (TRI) (7) has heightened the concern over the nation's air quality. Although this concern has been directed primarily at human health effects in urban-industrial areas, there is increasing concern among scientists that adverse ecological impacts may result from the deposition of toxic chemicals into natural ecosystems and the subsequent exposure of plants and other biota. The chronic exposure of vegetation to low concentrations of airborne toxic chemicals may result in sublethal effects, such as decreased plant productivity, vigor, and reproduction. Exposure may culminate in changes in plant community composition and ecosystem structure and function. This paper presents an overview of contaminant emission sources, atmospheric transport and deposition processes, evidence of the long-range transport of contaminants, and the potential effects of contaminants on terrestrial vegetation and ecosystems. Anthropogenic Emission Sources Although humans have been responsible for emitting contaminants into the atmosphere for thousands of years, air pollution has increased exponentially, both in quantity and variety, since the industrial revolution. Anthropogenic contaminants emanate from a host of different industrial, urban, and agricultural sources (Figure 1) such as: chemical, metal, plastic, and paper/pulp industries; fossil fuel processing plants; motor vehicles and aircraft; municipal waste incinerators; agricultural practices such as pesticide usage and field burning; and small businesses such as dry cleaners (7-9). Emissions of toxic chemicals into the atmosphere may occur directly, through deliberate or inadvertent release from industrial or urban sources, or indirectly, through volatilization following the deliberate or accidental discharge of chemicals into water or soil. Considerable amounts of toxic chemicals enter the atmosphere from wind drift and volatilization during and following agricultural pesticide applications (10). Glotfelty et al. (11) reported the significance of fog as an atmospheric phenomenon for concentrating and transporting pesticides at levels frequently exceeding 10 /*g/L.

Dunnette and O'Brien; The Science of Global Change ACS Symposium Series; American Chemical Society: Washington, DC, 1992.

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Contaminant Sources Point Sources CHEMICAL PLANTS METAL SMELTERS PULP & PAPER MILLS OR. REFINERIES POWER PLANTS WASTE INCINERATORS

Area Sources AGRICULTURE HOUSEHOLDS FORESTRY

Mobile Sources MOTOR VEHICLES AIRCRAFT

Biological Effects Contaminants

F o o d Chain Contamination

Industrial Organics PCBs HCB PCDOs PCDFs PAHs

Pesticides HCHs DDT TOXAPHENE CHLORDANES DIELDRIN

Abiotic Media

Bioaccumulation

H ORGANISM Altered Performance

ATRA2NE

SIMAZINE ALACHLOR

Trace Metals LEAD MERCURY CADMIUM ARSENIC ZINC NICKEL VANDIUM CHROMIUM

POPULATION O c c u r e n c e , A b u n d a n c e , Reproduction

COMMUNITY / ECOSYSTEM Structure, C o m p o s i t i o n , Function

Figure 1. Conceptual model illustrating examples of major anthropogenic contaminant sources and contaminants, their distribution within the abiotic environmental media, their movement into biota with potential food chain contamination, and potential effects at the organismal, population, community and ecosystem level of organization.


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Worldwide, over 63,000 chemicals are commonly used (12). The world's chemical industry markets an estimated 200 to 1,000 new synthetic chemicals, annually (13). Many of these chemicals eventually are emitted into the atmosphere. Industry is probably the major anthropogenic source of airborne toxic chemicals (7,14). According to the TRI estimates, United States industries emitted more than 1 χ 10 kg of toxic chemicals into the atmosphere, both in 1987 and 1988 (7). The TRI underestimated the actual air emissions as it did not include air emissions from numerous area sources (e.g., agriculture, households), mobile sources (e.g., motor vehicles), some industrial categories such as petroleum tank farms, federal facilities, companies with fewer than 10 employees, and urban businesses (e.g., dry cleaners), nor did the report consider volatilization of toxic chemicals from contaminated soils and water. Another group of environmental contaminants not considered by the TRI are the polycyclic aromatic hydrocarbons (PAHs), which are released into the atmosphere during the combustion of fossil fuels, waste incineration and agricultural burning (75). The application of pesticides to agricultural, forest and household lands is likely a significant source of atmospheric contaminants. Atmospheric loads of pesticide residues can arise as aerosols transported by wind during initial spraying, by volatilization from soil and plant surfaces, or by attachment to airborne soil particles. Agricultural lands account for approximately 75% of the pesticide usage in the United States (16). Approximately 4.55 χ 10 kg of pesticide active ingredients are used annually on 16% of the total land area of the United States (16). The magnitude of pesticide residues entering the atmosphere during and following application is not well known, but is likely significant (10). Aside from the obvious atmospheric contaminant loadings that occur during spray applications of pesticides, volatilization of deposited pesticides from soil and plant surfaces can be as large as 90% of the amount applied, even for chemicals with relatively low vapor pressures (17). In a regional study, Glotfelty et al. (18) reported that atmospheric transport and deposition resulted in low-level but widespread contamination of the Chesapeake Bay. Measurable concentrations of the herbicides, atrazine and simazine existed at all times of the year in the Maryland airshed. These authors estimated that annual pesticide deposition (summer rainfall only) into Chesapeake Bay during the early 1980s ranged from 0.6 to 1.2 metric tons of atrazine, 0.11 to 0.14 metric ton of simazine, 2.4 to 9.8 metric tons of alachlor, and 0.54 to 1.1 metric tons of toxaphene. Although numerous toxic chemicals are released from anthropogenic sources, organochlorine compounds and several trace metals are of particular concern. Organochlorines are significant environmental contaminants due to their high stability and persistence in the environment, their chronic toxicity, their proven ability for bioaccumulation and biomagnification in food chains, and the large quantities that have been manufactured, used, and released into environmental media (19-21). Organochlorines represent a large class of chemicals that includes synthetic industrial organics (and their by-products) such as polychlorinated biphenyls (PCBs), hexachlorobenzene (HCB), polychlorinated


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dibenzodioxins (PCDD), and polychlorinated dibenzofurans (PCDF), and pesticides such as DDT, hexachlorocyclohexane (HCH) and toxaphene. Unlike synthetic organic contaminants, airborne trace metals have significant natural sources such as volcanoes, wind-borne soil particles, sea-salt spray, forest fires, and various biogenic sources (22, 23). Global estimates of both natural and anthropogenic trace metal emissions into the atmosphere suggest, however, that urban-industrial sources contribute significantly to atmospheric trace metal inputs. For example, ratios of anthropogenic-to-natural emissions for lead, cadmium, vanadium, zinc, nickel, arsenic and mercury were reported to be approximately 27.7, 5.8, 3.1, 2.9, 1.9, 1.6, and 1.4, respectively (23). All trace metals, even those with essential biochemical functions, have the potential to produce adverse biological effects at excessive levels of exposure. However, trace metals such as mercury, cadmium, lead, and arsenic are of particular environmental concern because they are biologically nonessential and are toxic to most organisms at relatively low concentrations (24). The deposition of persistent synthetic organics and trace metals into terrestrial ecosystems not only results in increasing concentrations of these contaminants in vegetation and soils, but also increases the contamination and risk to organisms at higher trophic levels such as herbivores, detritivores, and carnivores (19, 20, 25, 26). Atmospheric Transport and Deposition Processes On a global scale, the atmosphere serves as the major pathway for the transport and deposition of contaminants from emission sources to terrestrial and aquatic ecosystem receptors (22, 27). Once a contaminant is airborne, the processes of atmospheric diffusion, transport, transformation, and deposition act to determine its fate. These processes are complex and the degree to which they influence the fate of a particular contaminant is dependent on its physico-chemical characteristics, the properties and concentrations of coexisting substances, and the prevailing meteorological conditions, including wind, precipitation, humidity, temperature, clouds, fog, and solar irradiation. The simultaneous atmospheric processes of diffusion and transport are responsible for the dispersion of contaminants after their initial release from emission sources (22). Gaseous and particulate contaminants are dispersed horizontally and vertically through the lower atmosphere by turbulent diffusion, vertical wind shear, and precipitation. Contaminant transport is a result of local, regional, and global air mass circulations. The atmospheric residence times of individual contaminants, along with the factors stated earlier, determine their transport distances. Depending on emission source factors and meteorological conditions, and on the their physical and chemical properties, airborne contaminants may be deposited close to the source or be carried great distances by the wind before being deposited to surface receptors. Atmospheric residence times depend upon such characteristics as mode and rate of emission, atmospheric transformations, physical state (gas, solid, or liquid), particle size, and chemical reactivity (9, 22, 28).



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Atmospheric aerosols (suspensions of solid or liquid particles in a gas) contain particles with diameters ranging from approximately 0.002/tm to 100 μτη (28). With respect to atmospheric chemistry, the most important particles are in the 0.002 μτη to 10 μτη range. Particles with diameters greater than 2.5 μτη are usually referred to as large or coarse particles, while those with diameters less than 2.5 μτη are identified as small or fine particles. Because of their relatively large size, coarse particles usually settle out of the atmosphere rapidly due to gravitational sedimentation. The smallest sized fraction (diameters less than 0.08 μτη) of the fine particle grouping, often referred to as Aitken nuclei, have short atmospheric lifetimes due to their rapid coagulation. The mid-sized fraction (diameters ranging between 0.08 μπι and 2 μτη) of the fine particle grouping, known as the accumulation mode, is considered significant for air pollutants as these particles contain high levels of organic and trace metal contaminants. Because of their small size, accumulation-mode, fine particles do not settle out of the atmosphere rapidly by gravitational sedimentation and are removed more slowly by dry and wet deposition (27). Consequently, fine particles in this size range tend to have longer atmospheric residence times, and the potential for long-range transport is greater. In general, short atmospheric residence times for contaminants correlate with coarse particle size, high reactivity (i.e., likely to be transformed to secondary products), and water solubility. Chemicals that remain as fine particles or that are sparingly water soluble may have atmospheric residence times of several weeks or months. Toxic chemicals that are persistent and have high vapor pressures are more likely to enter the atmosphere and reach remote areas. Many organochlorine compounds are transported over long distances because of their physico-chemical characteristics of relatively high volatility, low water solubility, and high chemical stability. Although high vapor pressure indicates greater partitioning of the chemical into the atmosphere, this factor alone cannot be used to discount the importance of the atmosphere as the transport mechanism of chemicals with low vapor pressures. For example, synthetic organics with low vapor pressures that also have low water solubilities tend to volatilize from water or moist soil surfaces into the atmosphere, despite their low vapor pressures (29, 30, 31, 32). Henry's law coefficients (ratio of vapor pressure to water solubility) is an important indicator of the significance of the atmospheric pathway for toxic organic contaminants (30, 31). In addition, many synthetic organics and trace metals are either emitted directly into the atmosphere as fine particles or are adsorbed on atmospheric particles. Retention and long-distance transport of fine particles by the atmosphere is considered significant. Transformation of parent contaminants into secondary products may occur during the processes of atmospheric diffusion and transport as a result of physical, chemical, and photochemical processes (22). Chemical conversion within the atmosphere may also change the physico-chemical characteristics of contaminants, dramatically altering their atmospheric residence times and fates from those of the parent contaminants. The complex reactions within the atmosphere that are driven by chemical processes such as hydroxyl scavenging


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or solar irradience may result in the formation of products that can be more or less toxic than the parent compounds. Deposition is the atmospheric removal process by which gaseous and particulate contaminants are transferred from the atmosphere to surface receptors - soil, vegetation, and surface waters (22, 27, 28, 32). This process has been conveniently separated into two categories - dry and wet deposition. Dry deposition is a direct transfer process that removes contaminants from the atmosphere without the intervention of precipitation, and therefore may occur continuously. Wet deposition involves the removal of contaminants from the atmosphere in an aqueous form and is therefore dependent on the precipitation events of rain, snow, or fog. Evidence of Long-Range Atmospheric Transport and Deposition The transport of airborne contaminants downwind from point sources has received a great deal of attention since the beginning of this century due to the damaging effects of the plumes on vegetation (33). Vegetation damage in areas surrounding pollutant point sources has generally decreased through emission control technologies, but adverse effects resulting from regionally distributed pollutants (e.g., oxidant air pollutants, acid precipitation precursors) still persist. During the last 10 to 20 years, however, the phenomenon of long-range atmospheric transport has drawn more attention and has been implicated in the wide distribution of anthropogenic contaminants on regional to global scales. Synthetic industrial organics, pesticide residues, and trace metals have been detected in the air, water, soil, and biota of rural and remote areas such as the Arctic and Subarctic (34-44), the Antarctic (45-47), high-elevation forests and lakes (48, 49), the Great Lakes (50, 51), peatlands, (52, 53, 54, 55), and open oceans and seas (56, 57, 58). Perhaps the best evidence of long-range atmospheric transport and deposition of contaminants is the data generated from investigations conducted in peatlands and arctic environments. Ombrotrophic peatland ecosystems are considered ideal for establishing trends in contaminant deposition (59). Ombrotrophic bogs are isolated from surface and ground waters, and thus receive all their hydrologie, nutrient, and mineral inputs from the atmosphere. Secondly, due to the acidity of bogs, microbial activity is low, resulting in reduced transformation and degradation of anthropogenic organic chemicals. Lastly, due to the bog's high organic matter content, hydrophobic contaminants adsorb strongly to peat, minimizing depositional mobility. Because of these attributes, dated peat cores have been used to reconstruct the historical record of environmental exposure of remote areas to atmospherically derived chemicals, such as synthetic organic contaminants, which have not been continuously measured at any site since the beginning of their commercial production and use. Using dated peat cores from ombrotrophic bogs, Rapaport and Eisenreich (53, 55) demonstrated unequivocal evidence for chronic atmospheric deposition of PCBs, DDT, HCHs, HCB, and toxaphene across the mid-latitudes of eastern North America, and correlated their historical accumulation rates with



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production and use in the United States. Although the production and use of PCBs, DDT, HCHs, and toxaphene have been banned or restricted in the United States, Rapaport and Eisenreich (55) concluded that atmospheric deposition of these organochlorines to peat bogs of eastern North America is still occurring, and that atmospherically derived fluxes of DDT to these peat bogs are approximately 10-20% of the levels that occurred during the peak DDT usage of the 1960s. They postulated that the recent flux of DDT is a result of long-range atmospheric transport from Mexico and Central America, where this pesticide is still used in substantial quantities (52). Arctic regions have few significant, local anthropogenic sources of contaminants. However, during the last decade, it has become increasingly evident that the Arctic is the receptor of long-range, atmospherically transported chemical contaminants originating from anthropogenic sources located in more southern latitudes. Synthetic industrial organics and pesticides such as PCBs, DDT, toxaphene, chlordane, HCB, HCHs, aldrin, and dieldrin, which are produced and used in urban-industrial and agricultural regions of temperate and subtropical latitudes of North America and Eurasia, have been detected in measurable quantities in the abiotic and biotic components of arctic ecosystems. For example, average air concentrations for two sites in the Canadian high Arctic during sampling periods in 1986,1987, and 1988 ranged between 183 and 577 pg/m for HCH, 74 and 189 pg/m for HCB, 35 and 44 pg/m for toxaphene, 15 and 38 pg/m for PCBs, 3 and 10 pg/m for chlordane, and 1 and 5 pg/m for DDT (ρ,ρ'-DDT + ρ,ρ'-DDE) (40, 43, 57). At three sites in the same geographic region, Gregor (42) reported that the annual snowpack concentration for total H C H in 1986 ranged between 650 and 11,106 pg/L. Larsson et al. (21) and Bidleman et al. (60) provide evidence of an atmospheric link for various organochlorine contaminants to arctic terrestrial and marine food chains, respectively. 3

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Environmental Partitioning and Vegetation Exposure Biota are exposed to toxic chemicals through the environmental media of air, water, and soil (Figure 1). After atmospheric deposition to terrestrial ecosystems, the fate of a contaminant depends on its environmental partitioning, which dictates its potential impact on vegetation and other biota (61). For example, trace metals tend to accumulate on soil surfaces by their adsorption to organic matter and clay particles (25). Trace metal accumulation may reduce plant growth and vigor through the disruption of nutrient uptake by the roots and decreased organic matter decomposition by soil microorganisms. Gaseous chemicals reside in the atmosphere with the potential to disrupt plant-leaf biochemical processes (e.g., photosynthesis, respiration) after absorption through the stomata or cuticle (32). Because of the lipophilic nature of many synthetic organics, the waxy cuticle of plant leaves may accumulate high levels of these substances (26, 62, 63). Transfer of toxic chemicals among ecosystem compartments often occurs. For example, trace metals may be absorbed by plant roots or deposited onto the


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leaves and then transferred to the soil through tissue loss and decay (64). Contaminants may also be passed along food chains through herbivory with the potential for biomagnification (19, 25, 63, 64). The deposition of airborne toxic chemicals deposited into agricultural ecosystems may contaminate human food resources (65).


Potential Impacts on Terrestrial Vegetation and Ecosystems Scientists have recognized that air pollutants such as ozone, sulfur dioxide, fluoride, acid precipitation, and certain trace metals can adversely impact agricultural and natural plant communities (61, 66-68). Emissions of sulfur dioxide, hydrogen fluoride, trace metals, and other toxics from pulp and paper mills, ore smelters, and power plants have severely reduced vegetation cover, biodiversity, and ecosystem integrity downwind from point sources (33, 61, 69, 70). In addition to the localized adverse effects near point sources, atmospheric pollutants have also caused regional damage to agricultural crops and natural plant communities through exposure to chemical oxidants such as ozone and peroxyacetyl nitrates, or acid precipitation (67, 68, 71, 72). Although the effects on vegetation from most criteria pollutants are well documented in the literature, little is known regarding the effects from airborne contaminants transported and deposited in rural and remote environments. Weinstein and Birk (67) suggest that the "chemical substances that may have the most substantial effect on terrestrial ecosystems over the long term are those that are dispersed over wide regions at concentrations that induce sub-lethal, chronic, physiological stress." These authors also suggest that changes in ecosystem structure and function from such chronic exposures may not be fully manifested for long periods, and once expressed these changes may be irreversible. The potential biological effects of airborne contaminants on terrestrial vegetation can be mediated through individual plants to the community and ecosystem (67). Although the adverse impacts cannot be specified in detail, as plant species and ecosystem types react differently to stress, chronic exposure to airborne contaminants may lead to a cascading effect in which the following stages may be observed (Figure 1): (1) disruption of biochemical or physiological processes of sensitive plant species resulting in altered performance (75), (2) reduction in growth, reproduction, and abundance of sensitive populations (74), and (3) alteration in the composition, structure, and function of plant communities and terrestrial ecosystems (25, 66, 75). The type and magnitude of these effects depends on the pattern of exposure (e.g., duration, concentration, frequency, season) that individual plants receive, their sensitivity to the contaminant, and the phytotoxicity of the chemical. This cascading effect may have been best demonstrated from interdisciplinary research addressing the consequences of chronic oxidant air pollution exposure to the mixed conifer forests of the San Bernardino Mountains of Southern California. Miller et al. (76) reported that chronic exposure to oxidant air pollutants resulted in decreased photosynthetic capacity, premature



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leaf fall, reduced growth and seed production, and lower nutritive content in the living foliage of sensitive pine species. Subsequently, the weakened trees became more susceptible to fungal disease and insect attack. Increased pine defoliation and mortality resulted in increased litter depth, hindering pine seedling establishment; while, encouraging oxidant pollution-tolerant, fire-adapted plant species establishment in the understory. Miller et al. (76) concluded that the gradual destruction of this pine-dominated forest will eventually result in a less desirable, self-perpetuating community of shrub and oak species that will inhibit the natural reestablishment of pine and other conifer species. After contaminant absorption by the plants through the leaves or roots, biochemical processes are the first affected. If enzymatic degradation detoxifies the pollutant, then no injury will occur. However, if enzymatic action cannot render the pollutant or its metabolites harmless, then alterations in plant metabolism may result in foliar injury, altered carbohydrate and nutrient allocation, and reduced growth and reproductive capability (72). The degree of impact to the plant depends on the toxicity of the pollutant and its exposure pattern. Acute exposures usually cause observable morphological damage, such as leaf lesions, stunted growth, or even death. Plant death resulting from acute exposure is usually localized when it does occur, for example, when an inordinate amount of toxic chemical exposure occurs via an accidental release or pesticide wind drift. Chronic, sublethal exposures may not induce observable morphological damage; they may, however, alter biochemical pathways, which can result in decreased vigor and productivity, altered phenology, loss of tissue, or reduced reproductive potential. Altered physiological processes cause a loss of vigor and render the plant more susceptible to insect damage or disease (74, 77). With continual exposure, even at sublethal concentrations, sensitive plant populations may decrease in numbers, allowing tolerant species to become dominant. Thus, shifts in plant community structure and composition could result in decreased biological diversity and altered ecosystem functions (74, 77). Plant damage resulting from acute air toxic exposures are usually limited in time and space as a result of control technology and legislation. However, sublethal, chronic exposure to airborne contaminants may predispose vegetation to other natural stressors and induce damage or mortality (77). Even though airborne contaminant damage may not cause permanent functional loss, the diversion of biochemical resources to repair the injury can inhibit normal plant functions and retard plant growth. Thus, physiological stress induced by airborne contaminants may predispose a plant to other stressors such as frost, drought, insects, or disease (74). When an airborne toxic chemical is introduced into a plant community, some plants will be more affected than others depending on individual tolerances endowed by their genotype, as well as on their phenology, and various modifying microclimatic variables. The sensitive plants or species that are no longer able to compete adequately with the tolerant plants or species will be partially or completely replaced. Some scientists propose that the widespread



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forest tree decline is not the result of a single agent but of an interaction among chronic exposures to air pollutants and natural stressors (78, 79). Airborne contaminants may also have indirect effects on vegetation by directly affecting other organisms critically associated with the plants. Soil microorganisms and invertebrates are critical in ecosystems for litter decomposition and nutrient cycling. Accumulation of trace metals within the organic horizon of the soil may limit organic matter decomposition and nutrient availability to plants (25). Many plants rely on insects for pollination. Airborne contaminants arising from anthropogenic activities (e.g., agricultural insecticide use, power plant emissions) have been shown to adversely impact beneficial insect populations (80, 81, 82), with the potential to result in inadequate flower pollination and subsequent seed and fruit set. The effects caused by airborne contaminants on vegetation can indirectly affect animals within the system through impacts on food chains and habitat requirements. The best documented effect is biomagnification of contaminants through the food chain (19, 83, 84). As vegetation provides substantial depositional surface area, and since plants are the beginning of the terrestrial food chains, contaminants accumulated by plants (either internally or as external foliar contamination) are made available to herbivores. Biomagnification of contaminants occurs when the organisms in the food chain do not have the ability to detoxify or eliminate the chemical from their systems, resulting in increased concentrations within the organism. Radio-ecological investigations of the lichen-caribou-man food chain convincingly demonstrated that radionuclide, particularly cesium-137 and strontium-90, concentrations increased through this relatively simple food chain and that radionuclide adsorption by aerial parts of plants was the most important entry route into the food chain (85, 86). In a study conducted on the Scandinavian peninsula, Larsson et al. (21) provides data demonstrating a positive correlation between the atmospheric deposition of PCBs, DDT, and lindane (7HCH) and the concentrations of these persistent contaminants contained in terrestrial herbivores and predators. The authors postulated that the entry route into the food chain was herbivory of contaminated vegetation. Biomagnification of contaminants through food chains has resulted in adverse consequences to animals, particularly carnivores (19). For example, the population decline of peregrine falcons in Great Britain during the 1950s and 1960s was caused by the contamination of their food chain by dieldrin (13). Potential impacts of contaminants on habitat are reductions in cover and quality. The loss of preferred habitat may leave animals more susceptible to prédation and disease. Loss of reproductive habitat may result in fewer animals reproducing in a given season or exposing the young to increased prédation. For some animal populations, then, habitat changes may lead to decreased reproduction, increased mortality, and increased emigration.


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Conclusion Numerous anthropogenic sources and activities are responsible for releasing a large volume of persistent and toxic chemicals into the atmosphere. As supported by scientific evidence, many of these contaminants are transported long distances and deposited in rural and remote locations. The impacts from the chronic deposition of airborne toxic chemicals on various levels of ecosystem organization and their potential interaction with natural stresses to induce antagonistic to synergistic effects are unknown. The fact that many airborne chemicals pose hazards to human health is only one aspect of the problem. The continued deposition of airborne toxic chemicals on a regional to global scale will affect public welfare if it results in adverse impacts on the structure and function of sensitive ecosystems. Acknowledgments The research described in this document has been funded wholly by the U.S. Environmental Protection Agency. This manuscript has been subjected to the Agency's peer and administrative review, and it has been approved for publication as an EPA document. Mention of trade names or commercial products does not constitute endorsement or recommendation for use. Literature Cited 1. 2. 3. 4. 5. 6. 7.

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Björseth, Α.; Lunde, G.; Lindskog, A. Atmos. Environ. 1979, 13, 45-53. Rahn, K.A. Atmos. Environ. 1981, 15, 1447-1455. Rahn, K.A.; Lowenthal, D.H. Science 1984, 223, 132-139. Jones, K.C.; Stratford, J.A.; Tidridge, P.; Waterhouse, K.S.; Johnston, A.E. Environ. Pollut. 1989, 56, 337-351. Atlas, E.L.; Schauffler, S. In Long Range Transport of Pesticides; Kurtz, D.A. Ed.; Lewis Publishers, Inc.: Chelsea, MI, 1990; pp 161-183. Levy, H., II. In Long Range Transport of Pesticides; Kurtz, D.A. Ed.; Lewis Publishers, Inc.: Chelsea, MI, 1990; pp 83-95. Toxics in the Community: National and Local Perspectives; U.S. Environmental Protection Agency: U.S. Government Printing Office, Washington, D.C., 1990; EPA560/4-90-017. Freedman, B.; Hutchinson, T.C. In Effect of Heavy Metal Pollution on Plants: Volume 2 Metals in the Environment; Lepp, N.W. Ed.; Applied Science Publishers: Englewood, NJ, 1981; pp 35-94. Schroeder, W.H.; Dobson, M.; Kane, D.M.; Johnson, N.D. JAPCA 1987, 37, 1267-1285. Waddel, T.E.; Bower, B.T. Managing Agricultural Chemicals in the Environment: the Case for a Multimedia Approach; The Conservation Foundation: Washington, D.C., 1988; pp 42-43. Glotfelty, D.E.; Seiber, J.N.; Liljedahl, L.A. Nature 1987, 325, 602-605. Maugh, T.H. Science 1978, 199, 162.


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